Background Organophosphate pesticides are heavily used in agriculture, and adverse associations with respiratory health in occupational settings have been reported. However, most of the evidence comes from studies where there were no biomarkers of exposure and no objective outcome measurement. Non-occupational chronic effects among residents living in agricultural communities are less well described.
Objective To evaluate associations between early-life organophosphate exposure and lung function of children living in an agricultural community.
Methods Participants were 279 children from the Center for the Health Assessment of Mothers and Children of Salinas (CHAMACOS) longitudinal birth cohort. The area under the curve for organophosphate exposure was determined by urinary diethyl and dimethyl dialkylphosphate metabolites of organophosphate pesticides, which were measured five times during childhood (6–60 months). Spirometry was performed at age 7 years. Regression models controlled for maternal smoking during pregnancy, season of birth, particulate matter concentrations with aerodynamic diameter ≤2.5 μm (PM2.5), breast feeding duration, mould and pets at home, distance of home from a highway, food insecurity, maternal education, season of spirometry, sex, height and technician.
Results Childhood diethyl, dimethyl and total dialkylphosphate concentrations were associated with significant decreases in lung function at age 7. Specifically, we found lower FEV1, (L/s) (ß=−0.16, 95% CI −0.30 to −0.02, p=0.03) and FVC (L) (ß=−0.17, 95% CI −0.34 to 0.01, p=0.06) per 10-fold increase of total dialkylphosphate levels.
Conclusions Early-life organophosphate exposure as assessed by dialkylphosphate concentrations was adversely associated with 7-year-old children's lung function.
- Paediatric Lung Disaese
Statistics from Altmetric.com
If you wish to reuse any or all of this article please use the link below which will take you to the Copyright Clearance Center’s RightsLink service. You will be able to get a quick price and instant permission to reuse the content in many different ways.
What is the key question?
Does prolonged early-life exposure to organophosphate pesticides (OPs), the most commonly used pesticide in agriculture, have an adverse effect on paediatric lung function?
What is the bottom line?
This study presents the first scientific evidence that non-occupational early-life exposure to OPs (ie, chronic low-level exposure to OPs at environmental relevant concentrations) is associated with decreased pulmonary function and may have a restrictive effect on children's lungs.
Why read on?
The causes for much paediatric respiratory disease are not fully understood; we present a new link between pesticides that are heavily used in agriculture and paediatric respiratory health that may be important to clinicians and researchers.
The aetiology of chronic paediatric respiratory disease, such as asthma, is not fully understood.1–3 Some environmental agents such as air pollution and tobacco smoke have been reported to be adversely associated with respiratory symptoms and impaired lung function,1 ,2 and others such as pesticides and household chemicals have been implicated.2 ,3
Although most residential uses of organophosphate pesticides (OPs) were phased out in the mid-2000s, they are still heavily applied in US agriculture with 15 million kilograms used in 2007 (36% of total insecticide use).4 ,5 This is reflected in the widespread detection of OP metabolites—dialkyl phosphate metabolites (DAPs)—in urine samples from the general US population.6
OPs can affect respiratory function by inhibition of acetylcholinesterase (AChE).7 Additionally, animal studies have reported that at doses below those that can cause AChE inhibition, OPs can induce airway hyper-reactivity.8
Occupational investigations have reported adverse associations between pesticides and respiratory health, including rhinitis, asthma, chronic bronchitis, cough and wheeze.9 ,10 A comparison of 89 pesticide sprayers with 25 controls found an inverse association between self-reported long-term pesticide exposure and forced expiratory flow at 25–75% (FEF25–75), and between short-term exposure as measured by serum cholinesterase and FEV1.11 Working for the agricultural sector was inversely associated with FEV1 (in ex-smokers) in 13 253 subjects in the European Community Respiratory Health Survey study.12 Reported occupational exposure to unspecified pesticides was inversely associated with FEV1 and FEV1/FVC in 11 851 subjects in the LifeLines cohort.13 A reduction of FEV1 and FVC was demonstrated among 25 Sri Lankan farmers occupationally exposed to OPs.14 In a non-occupational survey of 213 households in South Africa an adverse association between wheeze and use of insecticide in the home was reported,15 and in random household samples in rural Ethiopia, wheeze and the use of malathion (an OP pesticide) were associated.16
Reported paediatric respiratory symptoms were associated in a few studies with early-life, non-specific pesticide exposure in non-longitudinal designs.17 ,18 A study based on 14 065 participants aged ≤18 years from the National Health and Nutrition Examination Survey reported ambiguous results—an association between wheezing and dry cough and pesticide use in the kitchen and dining room, but no association with overall domestic use.19
We previously reported an association between respiratory symptoms at age 5 and 7 and early-life exposure to OP pesticides as assessed by urinary DAPs measured during pregnancy and childhood.20 These children were participants in the Center for the Health Assessment of Mothers and Children of Salinas (CHAMACOS) study, a longitudinal birth cohort investigating the health effects of environmental exposures on pregnant women and children living in the Salinas Valley, California.21 In this study, we examine the association of urinary DAP concentrations in pregnant women and their children in early childhood with spirometry at 7 years of age. Here we present the first report3 on an association between exposure to OP pesticides, as measured by DAPs and pulmonary lung function tests in children.
Study setting and design
Pregnant mothers were recruited to the CHAMACOS study during October 1999–October 2000. Women were eligible for the study if they were ≥18 years of age, at <20 weeks gestation and were planning to deliver at the county hospital, English or Spanish speaking and Medi-Cal (a state health insurance programme based on economic need) eligible.
Six hundred and one pregnant mothers were recruited to the cohort; 526 delivered live-born surviving singletons. Detailed methods are described elsewhere.21 Research protocols were approved by the University of California, Berkeley, Committee for the Protection of Human Subjects. Written informed consent was obtained from the mothers. Child assent was obtained at age 7.
We performed spirometry on 279 of these children at age 7. FEV1, FVC and FEF25–75 were available for 279, 250 and 250 children, respectively. Of the children for whom we obtained FEV1, FVC and FEF25–75, we had prenatal urinary DAPs for 275, 246 and 246 mothers and early childhood DAPs for 231, 206 and 206 children, respectively.
Information on covariates was obtained by maternal interviews, home visits conducted by trained personnel when the children were 6 and 12 months old and abstraction of prenatal and delivery records by a registered nurse. Mothers were also asked whether the child had been prescribed any medication for asthma or wheezing/whistling, or tightness in the chest. Women were interviewed twice during pregnancy (mean±SD=13.4±4.7, 26.5±2.6 weeks’ gestation), after delivery and when their children were 0.5, 1, 2, 3.5, 5 and 7 years old.
A clinical examination was performed when the child was 7, including maximum expiratory flow volume tests and height and weight measurements. Identical dry-seal spirometers were used in the study. Routine calibration was performed every morning. Tests were performed by bilingual and bicultural technicians specifically trained for the study. Three identical EasyOne spirometers were used by two technicians; 92% of the tests were performed by the same technician. Quality control was supervised by two physicians experienced in paediatric spirometry.
Each child performed a maximum of eight expiratory manoeuvres and up to three best acceptable tests were kept by the spirometric software. Each acceptable blow lasted at least 3 s. The children were coached to blow until the EasyOne signalled that the test had ended. All attempts were coached. Quality control was also achieved by verifying that the child did not lean forward; air did not leak out of the side; the child took enough air in and took a deep breath right from the beginning; blew enough air out; did not stop blowing too soon; and took a big smooth breath. All manoeuvres were reviewed again and verified by the two physicians to assure quality control. See online supplementary methods for more details.
Pesticide exposure: DAP metabolites
Six urinary DAP metabolites of OP pesticides comprised three diethyl (DEs: diethylphosphate, diethylthiophosphate and diethyldithiophosphate) and three dimethyl (DMs: dimethylphosphate, dimethylthiophosphate and dimethyldithiophosphate) phosphates were measured twice during pregnancy (M±SD=13.4±4.7 and 26.5±2.6 weeks, respectively) and five times during childhood when children were approximately 0.5, 1, 2, 3.5 and 5 years old. Maternal and child urine samples were stored at −80°C. Non-specific DAP metabolites were summed on a molar basis to calculate total DEs, total DMs and total DAPs.22 Analyses were conducted by the Division of Laboratory Science at the Centers for Disease Control and Prevention using gas chromatography-tandem mass spectrometry and quantified using isotope dilution calibration.23
For prenatal analysis, we examined diethyl phosphates (DEs), dimethyl phosphates (DMs) and total DAP concentrations (nmol/L) from maternal urinary samples collected at the first and second halves of pregnancy (0–20, 21–40 weeks’ gestation), as well as the average of these two measurements. For postnatal analysis, we calculated the area under the curve (AUC) from the five urinary metabolite measurements conducted during childhood using the trapezoidal method.20 For each time interval, we calculated the time-weighted average concentration by multiplication of time between measurements (years) by the average of the two measured concentrations. Time-weighted averages from each time interval were summed to calculate the AUC. Forty-three children were excluded from the AUC analysis owing to lack of DAP measurements at either 0.5 or 5 years, or lack of more than one measurement at ages 1, 2 and 3.5 years. If a child had only one missing DAP measurement at 1, 2, or 3.5 years (n=5), we imputed the mean of the two closest measures. DAP concentrations (in the first and second halves of pregnancy; the arithmetic average of the two pregnancy measurements; and the AUC of the childhood measurements) were log10 transformed. DAP concentrations were corrected for urinary dilution in maternal samples by dividing the DAP concentration by urinary specific gravity and in child samples by dividing by urinary creatinine.
We used general linear models (GLMs) to estimate the associations of prenatal and early childhood DAPs with FEV1, FVC, FEV1/FVC and FEF25–75. We estimated the associations between the highest spirometric measures for children who had one, two or three manoeuvres and for children who had at least two manoeuvres (ie, two or three manoeuvres). Covariates were selected based on directed acyclic graphs. We controlled for child's sex, height, child's age (months) and age squared, pets at home (at ages 5 and 7), household food insecurity score during the previous 12 months (at age 7; measured by using the US Household Food Security Instrument, Spanish version24), maternal education, season of spirometry (winter/spring/summer/autumn) and technician. We also controlled for covariates previously identified in our analysis of DAPs and respiratory symptoms20 (tables 3 and 4): maternal smoking during pregnancy, season of birth (mould/wet/pollen/dry), mean daily particulate matter concentrations with aerodynamic diameter ≤2.5 μm (PM2.5) during the first 3 months of life, breast feeding duration, signs of moderate/extensive mould at home visit (6 or 12 months) and distance (≤150 m) from a highway (6 or 12 months). Season of birth corresponds generally to other potential exposures that might play a causal role in respiratory disease (see online supplementary methods).
Potential selection bias due to exclusion from final models of children with missing outcome data or missing covariates was addressed by comparing our results with GLM models that included stabilised inverse probability weights25 ,26 (see online supplementary material).
We analysed the data using Stata (V.IC13.0; StataCorp, College Station, Texas, USA) for GLM models and R (V.2.14.2; R Foundation for Statistical Computing, Vienna, Austria) for Super Learner models. We set statistical significance at p<0.05 for all analyses. We defined borderline significance at 0.05<p<0.1.
Most cohort participants were born to Mexican immigrant mothers who had less than a high school education. Most mothers lived in a household with at least one farm worker and almost 40% reported food insecurity when the children were 7 years old (table 1). Mean±SD values of FEV1 (L/s), FVC (L), FEV1FVC ratio and FEF25–75 (L/s) were 1.70±0.46, 1.97±0.51, 0.89±0.06 and 2.29±0.82, respectively (table 2). The geometric means of specific gravity-adjusted total DAP, DE and DM concentrations during pregnancy were 145, 22 and 105 nmol/L, respectively. Child creatinine-adjusted total DAP concentrations decreased with age, averaging 229, 237, 214, 161 and 128 nmol/g creatinine at 0.5, 1, 2, 3.5 and 5 years of age, respectively (see online supplementary material and table E1).
Average DAP urinary concentrations in mothers during pregnancy were not significantly associated with lung function measurements (see online supplementary table E2). Estimates from models from the first and second half of pregnancy and from models that also included children who had only one lung function measurement were also non-significant (data not shown).
We found adverse associations, between the AUC of total DAPs, DEs and DMs concentrations measured in children's urine between 0.5 and 5 years old and FEV1, FVC and FEF25–75 measured at age 7 (table 3). Specifically, the highest FEV1 measured from children who had at least two acceptable manoeuvres was significantly associated with total DAPs (adjusted ß for a 10-fold increase in concentration (aß)=−0.16, 95% CI −0.30 to −0.02, p=0.03) and DEs ((aß)=−0.16, 95% CI −0.30 to −0.03, p=0.02) and borderline associated with DMs (aß=−0.12, 95% CI −0.25 to 0.02, p=0.08) (table 3). The highest FVC measured from children who had at least two acceptable manoeuvres was borderline associated with total DAPs (aß=−0.17, 95% CI −0.34 to 0.01, p=0.06) and DEs (aß=−0.17, 95% CI −0.33 to 0.00, p=0.06) and non-significantly associated with DMs (aß=−0.13, 95% CI −0.29 to 0.04, p=0.1) (table 3). Additionally, the highest FEF25–75 measured from children that had at least two acceptable manoeuvres was borderline associated with DEs (aß=−0.26, 95% CI −0.55 to 0.03, p=0.08) (table 3) and was not significantly associated with total DAPs or DMs. The FEV1/FVC ratio was not associated with any DAP measurement (table 4).
Similar results were obtained when we excluded children who had been prescribed medication for asthma, wheezing or tightness in the chest during the past 12 months and who had used any medication in the past 24 h before spirometry (see online supplementary tables E3, E6 and E7). Results were also similar when we included in the models children who had one, two or three acceptable manoeuvres and when we conducted minimally adjusted models (tables 3 and 4, see online supplementary tables E2–E7). Similar results were obtained when we did not adjust maternal DAP concentrations for specific gravity or child AUC levels for creatinine (data not shown). When we examined sex interactions in our models, we found no interaction by sex (p value for interaction: 0.3 to 0.6; data not shown). Estimates for both inverse probability weighted and unweighted regression models yielded similar results (data not shown), suggesting that selection bias did not substantially modify our results. The attributes of families included in this analysis (n=279) did not differ significantly from those of families not included, including urinary DAP concentrations during childhood, maternal asthma, maternal education, marital status, poverty category and child's birth weight. However, mothers of children included in this study were slightly older (mean age 26.5 vs 25.4, p=0.02) and breastfed the index child for longer (9.1 months vs 4.9, p<0.01) than those from the initial cohort (see online supplementary methods).
Although organophosphate pesticides are still widely used in modern agriculture,4 ,5 the effects of low-level exposure on lung function of residents living in agricultural communities have not been previously well studied.3 Our study provides the first evidence for an adverse association between exposure to OPs during childhood and pulmonary function of children. We assessed this relationship using a biomarker of exposure, urinary DAP metabolites, measured during the prenatal period and multiple times during childhood, in a prospective birth cohort design. Our findings support and extend the results of previous occupational studies of OP exposure and respiratory symptoms and function,3 case studies of paediatric OP poisonings27 and cross-sectional investigations of respiratory symptoms in adults and children following reported pesticide exposure.15–19 Our findings on pulmonary function support our previous analysis of an association between childhood DAPs and maternal report of child's respiratory symptoms,20 but unlike our previous study on symptoms, we found no association between in utero exposure and pulmonary function.
It is biologically plausible that chronic exposure to OPs might result in abnormalities of the lung. In contrast to the well-known acute respiratory effects of high-dose OP exposure, which include bronchoconstriction, pulmonary oedema and respiratory muscle paralysis,28 the chronic effects of low-dose OP exposure are less well understood. Recently, it has been reported that additional mechanisms, including inhibition of muscarinic receptors in the airways, may mediate effects of chronic exposure to OPs at environmental relevant concentrations—below those needed to inhibit AChE.8 However, more studies are needed to clarify the underlying mechanisms between chronic OP exposure and lung impairment.
Furthermore, because both FEV1 and FVC were associated with DAP levels, while the FEV1FVC ratio was not (0.3≤p≤0.9), we suggest that prolonged OP exposure may restrict the growth of lung function. Although some occupational studies have reported either a potentially obstructive29 or no effect30 of OP exposure, other studies suggest that a restrictive abnormality may be associated with occupational exposure to OPs.14 ,31 ,32 For example, Peiris-John et al14 reported an association of AChE levels between and during OP spraying seasons, and a reduction of FEV1 and FVC with a normal FEV1FVC ratio among 25 farmers occupationally exposed to OPs. However, our results for FVC and the FEV1FVC ratio should be interpreted with caution since collecting high-quality spirometric data function is particularly challenging in young children.33
Limitations of the study design include loss to follow-up and challenges in exposure assessment. Selection bias due to loss to follow-up is always a possible limitation in observational studies. However, the results of the sensitivity analysis we conducted imply that selection bias did not substantially modify our results. There are no long-term biomarkers of OP pesticide exposure. The available methods have several limitations, including a short half-life in the body, high variability in exposure and being class-specific rather than pesticide-specific.3 ,34 Owing to logistical challenges, we also used spot urine samples, which may be less representative of exposure than 24 h samples. However, we did previously find strong correlations between full-day 24 h samples and same-day spot samples.34 Finally, urinary DAPs may represent exposure to preformed metabolites in food or the environment and not direct exposure to parent compounds.35 Thus, our use of seven measurements collected from pregnancy to early childhood might have resulted in some exposure misclassification. Nevertheless, DAPs are commonly used in epidemiological investigations and they represent the current state-of-the-art method for assessing broad exposure to OPs,35 ,36 since there are few sensitive and specific assays for parent compounds in blood or pesticide-specific metabolites in urine. Moreover, any exposure misclassification, if it occurred, would have tended to bias our results towards the null hypothesis.
Strengths of our study include the prospective cohort design with a relatively large sample size; an objectively measured outcome, pulmonary function; and the use of a biomarker for OP exposure. Additionally, we used a biomarker that was measured twice in pregnancy and five times during early childhood, which allowed us to study the long-term effects that OPs might have on respiratory health. Moreover, the temporal sequence between OP exposure, measured during pregnancy and at ages 0.5–5 years of age and lung function, measured at age 7, allowed us to eliminate the potential for temporal bias.
In conclusion, our findings suggest that early-childhood exposure to OP pesticides is associated with decreased pulmonary function among school-age children living in an agricultural community in California. In our study, each 10-fold increase in concentrations of OP metabolites measured through early childhood (0.5–5 years of age) was associated with a 159 mL/s decrease in FEV1 in 7-year-old children. In comparison, 30 years ago, passive paediatric exposure to maternal cigarette smoke was found to be associated with a decrease in FEV1 of 101 mL/s after 5 years of exposure.1 Thus, this study adds exposure to OP pesticides to the growing list of environmental exposures, including air pollution, indoor cook stove smoke and environmental tobacco smoke,1 ,2 that may play a key role in the pathophysiology of chronic respiratory disease in children. We suggest that future studies should attempt to replicate our findings in different study populations and focus on the mechanisms by which OP exposure affects lung development and function. Given the widespread use of OP pesticides worldwide, we believe these findings deserve further attention.
We thank the CHAMACOS staff, students, community partners and participants and families, without whom this study would not have been possible. We especially thank Michelle Vedar, MPH, the CHAMACOS field office staff as well as Nina Holland, PhD and the staff of the UC Berkeley School of Public Health Biorepository for their assistance in specimen management, and Dana Barr, PhD and her staff at CDC for DAP measurements.
This web only file has been produced by the BMJ Publishing Group from an electronic file supplied by the author(s) and has not been edited for content.
- Data supplement 1 - Online supplement
Contributors RR: carried out the scientific literature search; analysed the data; prepared the tables; drafted the manuscript; BE, KGH and AB collected the data; RR, BE, JRB and KGH interpreted the data; BE, JRB, KGH, RBG, SM and AB provided critical revisions. All authors provided substantial contribution to the conception/design of work; approved the current version and state that it is ready to be published; and agree to be accountable for all aspects of the work in ensuring that questions related to the accuracy or integrity of any part of the work are appropriately investigated and resolved.
Funding This work was supported by the grants 2P01ES009605 from NIEHS and RD-82670901, RD-83171001 and RD-83451301 from the U.S. EPA (B.E., PI) and by a post-doctoral fellowship from the Environment and Health Fund (EHF), Jerusalem, Israel (RR). The contents of this article are solely the responsibility of the authors and do not necessarily represent the official views of the funders.
Competing interests AB has served as a consultant on cases unrelated to the topics covered in this paper and has participated as a member of the Board for The Organic Center, a non-profit organisation that provides information for scientific research about organic food and farming. JRB is the physician member of the California Air Resources Board, a paid position.
Patient consent Obtained.
Ethics approval Research protocols were approved by the University of California, Berkeley, Committee for the Protection of Human Subjects.
Provenance and peer review Not commissioned; externally peer reviewed.